AbstrAct

In this study, the contents of dust and associated heavy metals on roadside plants were investigated to assess their foliar transfer. The study was con­ducted at six different locations (four roadside and two industrial) near an industrial area in Bilaspur

(Chhattisgarh), India. Six metals (Fe, Mn, Pb, Cu, Cr, and Cd) were examined in this study. The con­centrations of heavy metals in foliar dust were found to be in the order of Fe>Mn>Pb>Cu>Cr>Cd. How­ever, this relative order changed in the case of leaf concentrations to Fe>Mn>Cd>Cu>Pb>Cr. The metal concentrations in the dust and leaves can be attributed mainly to industrial and vehicular emis­sions. In contrast to other metals, Cd showed signif­icant accumulation in the leaves compared to the re­spective dust samples. This study showed different patterns in the distributions of heavy metals between the dust deposited on the leaves and the metal accu­mulated in the leaves. These results suggest that the dust retention and heavy metal accumulation in na­tive plant species should be explored in an attempt to manage these hazardous metallic elements.

Key words: Toxic heavy metals, Accumulation, Urban roadsides, Phytomonitoring, Air Quality

1. INTRODUCTIONHazardous air pollutants (HAPs) are released from a

variety of manmade sources including industry, the combustion of fossil fuels, vehicular traffic (transport), and energy production. A large fraction of HAPs are “heavy metals” (Sawidis et al., 2011), including toxic trace elements such as Cu, Zn, Pd, Cd, and Cr. Vehicu-lar transportation is responsible for re-suspending and mixing fine particles in street dust (Zhang et al., 2012). Heavy metals in dust can exert direct effects on public

health because they can easily enter the human body via breathing, dermal contact, and dust ingestion, ulti-mately damaging the tissue of lungs (Zhang et al., 2012; Hu et al., 2011; Shi et al., 2011; Zheng et al., 2010; Ferreira et al., 2005; Drekert et al., 1991).

It has been reported that plants may be used as bio-logical filters by taking advantage of their foliar accu-mulation of particulate matter (PM) (Escobedo et al., 2008; Nowak et al., 2006). Plants can also be used as effective biomonitors to detect the presence of metals, even at trace levels, in the soil and in the atmosphere

(Sawidis et al., 2011). In recent years, a number of studies have reported the use of different plant parts as potential biomonitors of airborne heavy metals includ-ing (1) the leaves/needles of spruce (Brunner et al., 2008; Shparyk and Parpan, 2004), (2) birch (Kozlov, 2005), (3) pine (Przbysz et al., 2014; Serbula et al., 2013; Sawidis et al., 2011), (4) oak (Madejon et al., 2006), (5) olive (Madejon et al., 2006), (6) the bark of oak (Aboal et al., 2004), (7) pine (Patrick et al., 2007; Saarela et al., 2005), and (8) ash trees (Catinon et al., 2009). Hence, both leaves and bark can be used to monitor heavy metals (dust-bound) due to their high affinity for accumulation (Sawidis et al., 2011). Toma-sevic et al. (2005) described that the amount of PM deposited on leaves depends on the species and is re-lated to the different characteristics of the epidermis. Because most of these studies have been confined to developed regions around the world, there is a paucity of information from other regions, especially from India.

In this study, airborne heavy metals in dust particles that have been deposited on leaves were investigated to attain knowledge about the roadside contamination of hazardous air pollutants (HAPs) in Bilaspur. The present study seeks to quantify toxic heavy metals (in-cluding Pb, Cu, Cd, Mn, Fe, and Cr) in dust-deposited plant leaves and determine the extent of their uptake/accumulation in the leaves. Moreover, the dust-hold-ing capacities of different plant species were also cal-

Ozone Concentration in the Morning in Inland Kanto Region 137Asian Journal of Atmospheric EnvironmentVol. 10-3, pp. 137-145, September 2016doi: http://dx.doi.org/10.5572/ajae.2016.10.3.137

ISSN (Online) 2287-1160ISSN (Print) 1976-6912

Foliar transfer of Dust and Heavy Metals on roadside Plants in a subtropical Environment

Triratnesh Gajbhiye, Ki-Hyun Kim1),*, Sudhir Kumar Pandey* and Richard J. C. Brown2)

Department of Botany, Guru Ghasidas Central University, Bilaspur, 495009, C.G., India 1)Department of Civil & Environmental Engineering, Hanyang University, Seoul 04763, Republic of Korea 2)Environment Division, National Physical Laboratory, Teddington, Middlesex, TW11 0LW, UK

*Corresponding author. Tel: +91­7587194630, E­mail: skpbhu@gmail.com (S.K. Pandey) *Co­corresponding author. Tel: +82­2­2220­2325, E­mail: kkim61@hanyang.ac.kr (K.­H. Kim)

138 Asian Journal of Atmospheric Environment, Vol. 10(3), 137-145, 2016

culated to explore their possible role in dust nuisance management.

2. MaTeRIals aND MeThODs

2. 1 study areaBilaspur city is located in central India in the state of

Chhattisgarh. Its estimated population is 331030 with an area of 145.76 km2. This region is a semi-arid, sub-tropical zone. A map of the study area showing the study sites is presented in Fig. 1. Dust/plant samples were collected from six different locations (S1 to S6) along the roadside (Bilaspur to Sipat). Six plant species

(i.e., Mangifera indica, Pongamia pinnata, Calotropis procera, Kigelia pinnata, Butea monosperma, and Alstonia scholaris) were used for biomonitoring of dust-bound heavy metals. The first two sampling sites

(S1 and S2) were located inside the premises of the National Thermal Power Corporation (NTPC), which is a coal-based thermal power plant. The coal for the power plant is transported from the mines of South Eastern Coal Field Limited (SECL). Site 3 (S3) is located near the gate of the fly ash plant of the NTPC. The other three sites (S4 to S6) were roadside loca-tions with high traffic density (more than 3500 cars/heavy vehicles per hour). A detailed description of the selected sites is given in Table 1.

2. 2 sampling and sample PreparationPlant leaf samples were collected from all of the

study sites at a height of approximately 1.5 m (ambient height) in the month of January within a period of one day (January 28, 2014) to minimize temporal changes. These plants were selected because they are commonly

found throughout the city of Bilaspur. Samples were collected in Ziploc plastic bags and carried to the labo-ratory. Special care was taken to avoid loss of fine dust particles while separating dust from the sampled leaves. Dust was removed from the plants leaves and weighed. Leaf samples were washed, and their surface areas were calculated by a graph paper method. The leaves were oven dried for 24 h at 30°C and crushed into a fine powder. The weight of each sample (both dust and leaf powder samples) was approximately 2 g. Both dust and leaf powder samples were digested and pre-pared according to US EPA method 3050 B in order to analyze the heavy metals via atomic absorption spec-troscopy (US EPA 1996).

2. 3 analysis of MetalsAfter sample preparation, the heavy metal concentra-

tions of the samples were analyzed using flame atomic absorption spectroscopy (AA 7000, Shimadzu, Japan). The elements were measured against a 1000 μg mL-1 multi-element AA calibration standard solution (999±10 μg mL-1). A calibration curve was used to determine the concentrations of the elements. Blank corrections were also made from samples containing no dust. All concentrations are reported in μg g-1. The detection limits (DLs) of the six target metals were 0.04 μg g-1

(Fe), 0.01 μg g-1 (Mn), 0.08 μg g-1 (Cr), 0.08 μg g-1 (Pb), 0.006 μg g-1 (Cd), and 0.009 μg g-1 (Cu). The precision, when expressed as a relative standard deviation (RSD %), was below 5% for all of the metals.

2. 4 Dust-holding CapacityAfter cleaning, the collected leaves were put on graph

paper and outlined with a pencil. The leaf areas were calculated based on the graph squares. The dust-hold-

Fig. 1. Geographical map showing the sampling locations and study areas in Bilaspur (C.G.), India.

Foliar Transfer of Dust and Heavy Metals 139

ing capacities of the sampled leaves (from different sites) were calculated by the formula W/A (W = W2-W1)

whereW = total dust content (g)W2 = final weight of the paper with dustW1 = initial weight of the paperA = total area of leaf (cm2)

3. ResUlTs aND DIsCUssION

3. 1 Dust-holding Capacity of Different Plant species

As shown in Table 2, the highest dust-holding capa-city (g cm-2) was recorded for Calotropis procera

(0.0250). This was followed by Alstonia scholaris

(0.0042), Pongamia pinnata (0.0040), Mangifera indica

(0.0038), Kigelia pinnata (0.0030), and Butea mono-sperma (0.0025). Dust deposition and accumulation in different plant species can depend on a variety of fac-tors such as the leaf shape and size, orientation, tex-ture, presence/absence of hairs, and the length of the petioles. Higher dust deposition may be due to hairy, waxy coatings on the leaves with folded margins and rough surfaces. Lower depositions can be ascribed to the vertical position of the leaves. There was an in-verse correlation (r = -0.90, P>0.01, one-tailed) be-tween leaf area and the dust-holding capacity. This goes against the general expectation that a higher leaf area will hold more dust. In this work, it was found that instead of the leaf area (or leaf size), the plant type

Table 1. Description of the sampling sites.

Site No. Name of plants GPS location Site description Site pictures

S1 Mangifera indica N 22°07′19.2″ NTPC near the coal dump area. Coal particles are deposited everywhere.E 82°17′17.5″

S2 Pongamia pinnata N 22°07′09.4″ NTPC near the coal crushed house-II plant. Fine coal particles settled on plant parts.E 82°17′27.9″

S3 Calotropis procera N 22°08′11.4″ Near ash plant gate, heavy fly ash depositions on plants.E 82°17′05″

S4 Kigelia pinnata N 22°07′44.5″ Near a mandir, heavy traffic and industrial area.E 82°15′55.5″

S5 Butea monosperma N 22°07′13.9″ Near roadside, traffic area.E 82°14′31.8″

S6 Alstonia scholaris N 22°06′20.5″ Roadside, near rice mill, medium traffic.E 82°14′31.8″

140 Asian Journal of Atmospheric Environment, Vol. 10(3), 137-145, 2016

(species) is more important.

3. 2 Concentrations of Metals in Dust and leaves

The concentrations of heavy metals in the deposited dust and accumulated in the leaves are given in Table 3. The distribution behaviors of the individual metals that we measured are discussed below:Fe

Fe was found to be the dominant metal. In this study, the amount of Fe in the dust samples ranged from 1968

(at site 1) to 2103 μg g-1 (at site 3). Site 3 was near a fly ash dump area of the NTPC and had the highest density of heavy traffic (to transport the fly ash produced by the NTPC). The lowest Fe concentration was found at site 1; this is likely due to the fact that it had the lowest

level of traffic. However, in the case of the leaf sam-ples, site 5 (Butea monosperma) showed the highest accumulation of Fe (1669 μg g-1). Site 5 was situated near the roadside and had a high traffic load. At site 2, Pongamia pinnata had the lowest accumulation of Fe

(447 μg g-1).Mn

The amount of Mn in the dust samples ranged from 166 (at site 1) to 547 μg g-1 (at site 3). Due to the heavy traffic at site 3, Calotropis procera showed a high con-centration of Mn. There is a considerable difference in the Mn content between the different sampling sites. However, in the case of accumulation on the leaves, Butea monosperma recorded the highest concentration

(159 μg g-1) of Mn; this may be due to its larger sur-face. The lowest concentration of Mn was observed at site 6 (Alstonia scholaris).Cr

The Cr concentration in the dust ranged from 6.60

(at site 1) to 30.6 μg g-1 (at site 3). At site 3, a large amount of fly ash dust was deposited on plant leaves near the fly ash plant of the NTPC. Moreover, this site is also affected by a heavy traffic load. The amount of Cr in the dust can be affected by the chrome plating of some motor vehicle parts (Alshayep and Seaward, 2001). The lowest level of Cr was found at site 1, where very little traffic activity was observed. Among the leaves, the highest concentration of Cr (27.9 μg g-1)

Table 3.

(a) Concentrations of metals deposited on leaf surfaces in the dust (μg g-1).

S. No. MetalS1 S2 S3 S4 S5 S6

Mangifera indicia

Pongamia pinnata

Calotropis procera

Kigelia pinnata

Butea monosperma

Alstonia scholaris

1 Fe 1968 2014 2103 2100 2086 20992 Mn 166 183 547 473 455 5293 Cr 6.60 7.80 30.6 16.5 14.4 15.04 Pb 9.18 27.9 24.8 16.5 25.7 23.65 Cd 0.06 0.63 0.09 1.31 0.38 0.546 Cu 12.5 8.11 17.1 27.7 22.9 21.1

(b) Concentrations of metals accumulated in the leaves (μg g-1).

S. No. MetalS1 S2 S3 S4 S5 S6

Mangifera indica

Pongamia pinnata

Calotropis procera

Kigelia pinnata

Butea monosperma

Alstonia scholaris

1 Fe 447 301 1080 1294 1669 7162 Mn 158 130 143 64.9 159 45.83 Cr 27.9 2.10 7.20 3.60 3.30 1.804 Pb 1.22 11.9 11.6 12.6 11.3 11.95 Cd 13.6 14.5 13.7 13.0 12.3 11.86 Cu 27.5 8.89 5.63 9.33 11.2 3.50

Table 2. Dust-holding capacity (DHC) calculated for differ-ent plant species at different sites (Dust weight for all of the samples was 2 g).

Site Plant species Leaf area (cm2) DHC (g cm-2)

S1 Mangifera indica 520 0.0038S2 Pongamia pinnata 502 0.0040S3 Calotropis procera 80 0.0250S4 Kigelia pinnata 660 0.0030S5 Butea monosperma 794 0.0025S6 Alstonia scholaris 476 0.0042

Foliar Transfer of Dust and Heavy Metals 141

was observed at site 1 (Mangifera indica). This was situated in a coal dump area. The lowest Cr concentra-tion was found at site 6 (Alstonia scholaris).Pb

The Pb concentration in the dust ranged from 9.18

(at site 1) to 27.9 μg g-1 (at site 2). Concentrations of Pb in the deposited dust samples were reported to be mainly caused by the traffic activity due to the utiliza-tion of leaded gasoline (Day et al., 1975; Yongming et al., 2006). The other sampling sites showed a range of concentrations, indicating the variable levels of vehic-ular activities.

In the leaves, the highest Pb value (12.6 μg g-1) was found at site 4 (Kigelia pinnata). This site was near a road junction with heavy traffic. Hence, the large amount of leaded petrol emissions on the leaves of Kigelia pinnata at this location likely contributed to the highest accumulation of Pb. Site 1 (Mangifera indica) had the lowest Pb accumulation (1.22 μg g-1) because it was located at a coal dump area with negli-gible traffic.Cd

In the case of the dust samples, the concentration of Cd ranged from 0.09 (at site 3) to 1.31 μg g-1 (at site 4). Interestingly, it was below the detection limit (0.006

μg g-1) at site 1. The concentration of Cd in the leaves showed the highest value at site 2 in Pongamia pinnata

(14.5 μg g-1). If we compare the concentration values of Cd in the dust against those in the leaves, its ratio ranged from 10 (in leaves of Kigelia pinnata at site 4) to more than 100 (in leaves of Calotropis procera at site 3). Hence, it appears that Cd was the most accumulat-ed toxic metal in plant leaves (from dust and/or other sources, mostly airborne) at all of the sites. Calotropis procera showed the highest accumulation potential for foliar uptake of Cd.Cu

The concentration of copper in the dust ranged be-tween 8.11 (at site 2) to 27.7 μg g-1 (at site 4). The source of copper in street dust can be attributed to the abrasion of metallic parts of vehicles caused by engine

wear, brushing, and bearing metals (Al-khashman and Shawabkeh, 2006; Al-Khashman, 2004). Interestingly, at site 4, there was a speed bump; copper can be re-leased from brake linings as vehicles stop and start. At site 1, Mangifera indica showed the highest concentra-tion of Cu (27.5 μg g-1) among the leaves. The mini-mum value of Cu in the leaves was 3.50 μg g-1 at site 6

(Alstonia scholaris). The relatively high concentration of Cu in these leaves showed the high accumulation potential of Mangifera indica.

3. 3 Overall Distribution Pattern of Target heavy Metals

In order to obtain an overall picture of the distribu-tions and relative contributions of the different metals, the mean concentration values of each metal were com-puted from the different sites (Table 4). As shown in Table 4, Fe constituted the major fraction among all of the target metals, showing a concentration of 2062±56.8 μg g-1. This was followed by Mn (392±172 μg

g-1), Pb (21.3±7.06 μg g-1), Cu (18.2±7.16 μg g-1), Cr

(15.2±8.58 μg g-1), and Cd (0.48±0.50 μg g-1). How-ever, in the leaves, the order changed to Fe>Mn>Cd >Cu>Pb>Cr. Moreover, all of the metals showed significantly positive correlations between the dust concentrations and the leaf concentrations, suggesting that a certain fraction of the metals are transferred from the dust to the leaves (Table 5). Hence, if we assume that all of these toxic metals are due to the airborne dust that is released from vehicular and industrial sources, the accumulation of toxic metals should depend on the location relative to the emission sources. Additionally, the leaf concentrations varied across different plants at different sites in the order of Butea monosperma> Calotropis procera>Kigelia pinnata> Alstonia scholaris>Mangifera indica>Pongamia pinnata. This may reflect variations in both plant characteristics and source-related activities.

3. 4 Factors affecting the Distribution Behavior of heavy Metals

A correlation analysis was performed between the

Table 4. Statistical parameters for the distribution of target heavy metals in the dust deposited on the leaves and in the leaves from the selected study areas.

Metal Fe Mn Cr Pb Cd Cu

All site

(Leaf dust)Mean±SD 2062±56.8 392±172 15.2±8.58 21.3±7.06 0.48±0.50 18.2±7.16Min-Max

(Median)1968-2103

(2093)166-547

(464)6.60-30.6

(14.7)9.18-27.86

(24.2)0-1.31

(0.46)8.11-27.7

(19.1)

All site

(Leaves)Mean±SD 918±524 117±49.1 7.65±10.1 10.1±4.37 13.2±0.99 11.0±8.54Min-Max

(Median)301-1669

(898)45.8-159

(137)1.80-27.9

(3.45)1.22-12.6

(11.8)11.8-14.5

(13.3)3.50-27.5

(9.11)

142 Asian Journal of Atmospheric Environment, Vol. 10(3), 137-145, 2016

different metals (Table 6). According to the correlation analysis, there were significant positive correlations between pairs of Mn/Fe (r = 0.97, P<0.01), Cr/Mn

(r = 0.80, P<0.05), Cu/Fe (r = 0.76, P<0.05), Cu/Mn

(r = 0.76, P<0.05), and Fe/Cr (r = 0.74, P<0.05). This observation indicates that dust contamination by metals may originate from common anthropogenic sources.

Mn and Fe are the most dominant metals in the depos-ited dust. It was noted that, other than the NTPC, there is no heavy (or major) industrial development near the sampling sites; thus, the target heavy metals in the deposited dust appear to be derived mainly from auto-mobiles.

In the leaves, Pb/Cr (r = -0.98, P<0.01) and Pb/Cu

(r = -0.94, P<0.01) consistently showed inverse cor-relations. Such a strong inverse correlation between Pb and Cr suggests their competing potential for uptake/accumulation. In addition, Cr/Cu showed a strong pos-itive correlation (r = 0.92, P<0.01).

Statistical analysis revealed that some metals are strongly accumulated by specific plants. For instance, in the case of Fe, Mangifera indica, Calotropis procera, and Kigelia pinnata showed a strong correlation be-tween the dust and leaf concentrations. Hence, Man-gifera indica, Calotropis procera, and Kigelia pinnata are shown to be efficient accumulators of Fe. Similarly, in the case of Mn, Mangifera indica, Pongamia pinna-ta, Kigelia pinnata, and Alstonia scholaris showed significant accumulation. For Cr, Pongamia pinnata, Calotropis procera, Kigelia pinnata, and Butea mono-sperma were found to be good accumulators. For Pb, Mangifera indica, Pongamia pinnata, Calotropis proc-era, and Butea monosperma were good accumulators. For Cd, Mangifera indica, Calotropis procera, and Kigelia pinnata showed good performance in terms of metal accumulation. For Cu, Mangifera indica, Kigelia pinnata, and Butea monosperma showed a superior correlation coefficient. Moreover, it is important to note that Mn, Cr, and Pb showed good correlations (P<0.01 level), suggesting that these metals are heavily accu-mulated in these plants (Table 7).

3. 5 Comparison between Different studiesThe concentrations of heavy metals reported in pre-

vious studies (deposited dust samples and/or leaf accu-mulation) are compared with this study in Table 8. The coal-based thermal plant and roadside traffic activities should be the main sources of heavy metal pollution at the study site. In Calcutta, India, the concentrations of

Table 5. Correlation of metals between leaves and dust across different sites (plants).

Plants Correlation (r) Metals

Mangifera indica 0.96** Fe, Mn, Cr, Pb, Cd, CuPongamia pinnata 0.95** Fe, Mn, Cr, Pb, Cd, CuCalotropis procera 0.99** Fe, Mn, Cr, Pb, Cd, CuKigelia pinnata 0.98** Fe, Mn, Cr, Pb, Cd, CuButea monosperma 0.99** Fe, Mn, Cr, Pb, Cd, CuAlstonia scholaris 0.98** Fe, Mn, Cr, Pb, Cd, Cu

**Correlation is significant at 0.01 level (one-tailed)

Table 6. Results of correlation analysis: Factors affecting the distribution of heavy metals.

(a) Dust on leaves

Fe Mn Cr Pb Cd Cu

Fe 1Mn 0.97** 1Cr 0.74* 0.80* 1Pb 0.49 0.35 0.33 1Cd 0.45 0.26 -0.04 0.15 1Cu 0.76* 0.76* 0.37 -0.07 0.56 1

(b) Leaves

Fe Mn Cr Pb Cd Cu

Fe 1Mn 0.02 1Cr -0.37 0.48 1Pb 0.42 -0.48 -0.98** 1Cd -0.53 0.49 0.27 -0.21 1Cu -0.28 0.54 0.92** -0.94** 0.28 1

*Correlation is significant at 0.05 level (one-tailed)**Correlation is significant at 0.01 level (one-tailed)

Table 7. Correlation of metals between leaves and dust in selected plants of all the sites.

Metal Correlation (r) Plants considered (showed the best correlation results)

Fe 0.96 Mangifera indica, Calotropis procera, Kigelia pinnataMn 0.98** Mangifera indica, Pongamia pinnata, Kigelia pinnata, Alstonia scholarisCr 0.995** Pongamia pinnata, Calotropis procera, Kigelia pinnata, Butea monospermaPb 0.99** Mangifera indica, Pongamia pinnata, Calotropis procera, Butea monospermaCd 0.97 Mangifera indica, Calotropis procera, Kigelia pinnataCu 0.98 Mangifera indica, Kigelia pinnata, Butea monosperma

*Correlation is significant at 0.05 level (one-tailed)**Correlation is significant at 0.01 level (one-tailed)

Foliar Transfer of Dust and Heavy Metals 143

metals (Fe, Mn, and Pb) were the highest in both de-posited dust and leaf samples, where the main sources were heavy traffic activities, industrial emissions (such as a Pb factory), and the use of agricultural chemicals. In the deposited dust, the mean Fe concentration of the present study (2061 μg g-1) was considerably lower than that of Calcutta (21800 μg g-1); the Fe concentra-tions in this study were roughly one order of magnitude lower than those in Calcutta. Alternatively, the mean concentration of Mn (329 μg g-1) in the deposited dust was nearly 2.5 times lower than that of Calcutta (820

μg g-1) and two times lower than that of Hangzhou

(526.7 μg g-1). In the case of Hangzhou, the major sources of heavy metals were suggested to be coal com-bustion, traffic emissions, and industrial activity.

The mean levels of Cr (15.2 μg g-1) in the deposited dust of Bilaspur were much lower than those of other cities; these values were six times lower than Calcutta

(97 μg g-1), five times lower than Hangzhou (73.3 μg

g-1), and 24 times lower than Huizhou (364 μg g-1). The highest concentrations of Cd and Pb were report-ed at Huizhaou; these were caused by the combined effects of many strong sources such as industrial, com-mercial, and traffic activities. The lowest value of Fe was reported in Calcutta (2.18 μg g-1) which was near-ly three orders of magnitude lower than the concentra-tion reported in our study. Alternatively, the mean con-centration of Mn (329 μg g-1) in our deposited dust was nearly 2.5 times lower than Calcutta (820 μg g-1) and two times lower than Hangzhou (526.7 μg g-1). The mean level of Cr (15.2 μg g-1) in the deposited dust of Bilaspur was almost six times lower than Cal-cutta (97 μg g-1), five times lower than Hangzhou (73.3

μg g-1), and 24 times lower than Huizhou (364 μg g-1). Similarly, the Pb (21.3 μg g-1), Cd (0.48 μg g-1), and Cu (18.2 μg g-1) concentrations in our study were pres-ent at lower levels than were reported in the literature.

In the leaf samples, the concentration of Fe in our study was 918 μg g-1, which was 41 times lower than Calcutta (3800 μg g-1). However, it was 2.5 and four times higher than the West Bank (349 μg g-1) and the city of Huelva (233.1 μg g-1), respectively. The accu-mulation of Mn (117 μg g-1) in Bilaspur (the present study) is nearly 1.5 times higher than that of the West Bank (71.8 μg g-1), which has high traffic activity. In contrast, it was 3.4 times higher than that of Huelva

(35.45 μg g-1), which is subject to industrial emissions. Finally, it was 1.2 times lower than that of Calcutta

(141 μg g-1), which is affected mostly by traffic and industrial sources.

In the leaves, the concentration of Fe in this study was 918 μg g-1, which was more than three orders of magnitude higher than Calcutta (0.38 μg g-1), 2.5 times higher than the West Bank (349 μg g-1), and four times higher than the city of Huelva (233.1 μg g-1). The ac-cumulation of Mn (117 μg g-1) in Bilaspur (the present study) was nearly 1.5 times higher than the West Bank

(71.8 μg g-1), 3.4 times higher than Huelva (35.45 μg

g-1), and approximately 1.2 times lower than Calcutta

(141 μg g-1). Similar results were found for Cr (7.65 μg

g-1) and Pb (10.1 μg g-1). However, the levels of Cu

(11 μg g-1) in this study were generally lower than pre-viously reported results (Table 8). Cd concentrations in the leaf samples in this study were more than two or-ders of magnitude higher than both Calcutta (0.47 μg

g-1) and the West Bank (0.14 μg g-1). Hence, the trans-fer of heavy metals from deposited dust to plant leaves appears to be governed by the combined effects of the type of plant and the type of metal.

4. CONClUsIONIn this study, six heavy metals (Fe, Mn, Cr, Pb, Cd,

Table 8. Comparison with previous studies or standards (all concentrations are in μg g-1).

(a) Dust deposited on leaves

City Fe Mn Cr Pb Cd Cu Reference

Calcutta 2.18 (%) 21800 820 97 1030 1.78 269 Chatterjee and Banerjee (1999)Hangzhou 45.6 526.7 73.3 150.9 2.62 63.7 Lu et al. (2008)Huizhou - - 364.7 410.4 8.6 603.3 Qiu et al. (2009)Bilaspur 2061 392 15.2 21.3 0.48 18.2 Present Study

(b) Metal accumulated in leaves

City Fe Mn Cr Pb Cd Cu Reference

Calcutta 0.38 (%) 3800 141 16.6 214 0.47 40 Chatterjee and Banerjee (1999)West bank 349 71.8 2.63 1.40 0.14 14.5 Swaileh et al. (2004)Huelva city 233.1 35.45 0.43 2.85 - 24.15 Oliva and Mingorance (2006)Bilaspur 918 117 7.65 10.1 13.2 11 Present Study

144 Asian Journal of Atmospheric Environment, Vol. 10(3), 137-145, 2016

and Cu) were investigated in dust samples with respect to their possible transfer and uptake in plant leaves. If we compare specific metal concentrations, Fe is domi-nant compared to all of the other metals in both the dust and leaf samples. Cd showed the highest accumu-lation potential in plant leaves from the dust compared to the other metals. Calotropis procera showed the highest accumulation potential for Cd. The significant inverse correlation found between the leaf area and the dust-holding capacity revealed that, instead of the leaf area (or leaf size), the plant type (species) is the most important factor. Hence, the plants growing in affected areas should be investigated for their metal accumula-tion potential in order to use them for possible moni-toring of toxic species in air.

aCkNOwleDgeMeNTThe first author is thankful for financial support from

the UGC, New Delhi, India for Rajiv Gandhi National Fellowship (RGNF). The corresponding author acknow-ledges financial support from a UGC start-up grant, New Delhi, India (No.F. 20-1/2012(BSR)/20-2(3)/2012 (BSR)) and a UGC-MRP grant (F. No.-43-311/2014

(SR)). The second author is thankful for a grant sup-ported from the National Research Foundation of Korea

(NRF) funded by the Ministry of Education, Science, and Technology (MEST) (No. 2006-0093848).

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(Received 13 May 2016, revised 3 August 2016, accepted 8 September 2016)